Treatment of fly ash from coal combustion to improve its marketability

ABSTRACT

A system and method for treating unmarketable fly ash and improve its properties as an additive for concrete is disclosed. The method includes the steps of providing a gas stream containing ionized air ( 34 ), and an amount of fly ash ( 10 ) containing carbon having an adsorption capacity. The fly ash ( 10 ) is then exposed to the gas stream ( 34 ) to expose the carbon to the ionized air to promote the attachment of the ions to the carbon to reduce the adsorption capacity of the carbon.

TECHNICAL FIELD

Coal combustion fly ash has been marketed for a variety of applications. The addition of fly ash to cement is an expanding industry and accounts for a huge opportunity for the coal burning power plants to defray operating costs for disposal. However if the ash does not meet certain guidelines in terms of residual carbon; or has surfactant adsorption problems-measured in terms of a foam index; or contains ammonia, the fly ash is not only unusable but becomes a disposal problem. This application is concerned with ways and means to treat unmarketable fly ash and improve its properties, use and value. It is of great importance to the power, cement and construction industries.

BACKGROUND ART

Fly ash derived from power plants is frequently used in the production of concrete. According to the relevant ASTM requirements, fly ash may replace cement in concrete up to 5-10%. Generally speaking if the carbon in the fly ash were less than 3% w/w (usually measured as loss in ignition or LOI, which closely correlates with the carbon content) it would be marketable. This is common with the C class ashes, which are generally from sub-bituminous coals. Quite often the bituminous coals, which lead to F class ashes, have much higher carbon levels and may in any event be unmarketable unless the carbon is burned out or removed by a separation process.

In the preparation of concrete known as “ready mix” air-entraining agents are used to allow the introduction of micro bubbles into the concrete. These micro bubbles aid in the control of expansion and contraction of the concrete as occurs with freeze and thaw in the environment. Too much air entrained in the concrete reduces strength and too little results in poor adaptation to the above weathering impacts. Many of the ashes can have a seemingly low carbon or LOI level and yet have a problem with the quantity of surfactant required to entrain micro bubbles. It has been determined that it is the carbonaceous residual in fly ash impacts the adsorption of surfactants. This carbon has a high surface area and is very active towards the so-called air entraining agents.

The normal cause of the problem with the fly ash is: low and ultra low NOx burner systems starve the combustion of the coal in the primary firing zone and then add over-fire air to complete oxidation. While minimizing NOx formation these conditions can create higher levels of condensed organic carbonaceous intermediates or soot in or on the fly ash, as well as incompletely combusted particles of (devolatilized) coal. They are effectively incomplete combustion products of the carbon. The remaining mineral matter then has a significant quantity of both coarse (−50 microns) and nano-particulate carbon intermingled with it.

-   -   This material has a tendency to adsorb the surfactants or air         entraining agents causing a high “foam index” and it is thought         that it is the finer particles that create most of the problem.         This high foam index relates to the number of drops of a         standard surfactant that is added to a known quantity of fly ash         under controlled conditions. A high foam index material requires         much more surfactant than normally necessary.

It is not often clear whether the cause of the high foam index is the reducing conditions in the combustion zone, the residence time of solids in the gas phase, or the load on the boiler unit. It is most probably a function of the specific surface area per unit volume of the carbon, which is related inversely to the particle size (diameter). These effects are not fully understood. Suffice it to say, there are many plants that have this problem with their fly ash. They are struggling to find a solution to overcome the issue so the ash may be sold rather than disposed. Additionally, the situation is worsened by the lack of knowledge of the correlation with the potential causes and the variability of the foam index value. It will be clear to the reader that the variable nature of the foam index will lead to an unknown or un-quantifiable amount of air entraining agent—one minute the amount added if constant might be too much and the next too little.

Another problem with fly ash arises from the presence of ammonia. If too high a concentration is present in the fly ash it may release upon addition of water and the other cement components leading to deleterious environmental consequences. Emission of ammonia is not only unpleasant in closed-in working environments; it is also toxic in high enough concentrations.

Ammonia in fly ash from power plants is created by the injection of ammonia to remove NOx. This technique is employed with Selective Catalytic Reduction (SCR) units. These control devices employ special catalysts, which combine ammonia with NOx components and form harmless nitrogen and water. Some stoichiometric excess is needed to assure the removal of the NOx, but over-injection creates ammonia “slip”, as it is referred to, which results in high local concentrations of the undesirable component adsorbed onto the particulates (or fly ash) in the gas stream. A′material so affected is difficult to sell into the concrete market.

These two problems occur in fly ash resulting from coal burning power plants where there are emission control features installed on the boilers. There are innumerable cases where there is need for correction of the either of II) the two issues and sometimes both on the same plant.

Thermal oxidation is a process that can remove both the ammonia and the carbon foam index issue. Indeed, carbon burn out facilities have been constructed that will take the carbon content and burn it to a low level and it is known that the foam index problem is destroyed under these circumstances. Temperatures for such processes are generally in the region of 700-850° C. Ammonia is also broken down by thermal oxidation means and this can take place at lower temperatures around 350 to 500° C.

Where the foam index issue has to be addressed without real burnout of the carbon (usually because there is insufficient to provide combustible heat release of any magnitude) the foam index can be ameliorated or lessened by thermal treatment at temperatures as low as 400° C. but generally more like 700° C. Naturally the requirement to heat up the fly ash to any of these temperatures results in the expenditure of quite a lot of energy or fuel. Some of this can of course be recovered in the gas stream to preheat the feed air for the combustion process, but nevertheless the demand for fuel is quite significant.

For the treatment of foam index problems, Hurt et al U.S. Pat. Nos. 6,136,089 and 6,521,037 have proposed and patented the use of ozone. This has the advantage of being applied at low temperatures negating the fuel requirements of a truly thermal or combustion process. The dosage rates are relatively high, though, and the use of ozone has an energy demand of its own. First, the production of ozone is inefficient due to side reactions and the overall power required for a reasonable concentration is quite significant. Secondly, ozone is made from an air stream or an oxygen stream or a mixture of both—but the gas must be almost completely dry (free of water). The generally known conditions for its production are a low dew point of −40° C. or lower in the gas stream, as it is unstable in moist air. Hence, an important part of the power consumed in its generation comes from the drying of the air stream to low dew points. Alternatively, oxygen may be used (which has an inherently low dew point due to the manufacturing processes—from cryogenics or pressure swing methods both of which eliminate water from the gas as an early step in the process chain). However, the power for production of oxygen has to be taken into account—this can range from about 200-400 kWh/ton. Oxygen enables higher concentrations of ozone to be made. Ozone made from oxygen can, for example, be as high as 1-6% w/w. Whereas the concentration level is significantly lower with air perhaps 200 ppm to 5,000 or 10,000 ppm.

The reaction, which produces ozone from a corona discharge in air or oxygen, is quite endothermic. The inefficiencies in the process lead to the release of energy as heat. This heat must be removed from the gas during production. If this heat is not removed, by a cooling circuit, the ozone breaks down—and effectively the product concentration is lowered significantly. The cost associated with the cooling duty is an additional power load and is often not figured in the production cost of ozone generators. This is the third source of cost.

Lastly, the capital cost of ozone generators is significant, as they require close tolerance in manufacture for fitting the dielectric inserts and electrodes within the tubular arrays in a concentric manner. This impacts the overall operating cost in terms of depreciation charges.

The power associated with production is in the range of 9 to 18 kWh/kg of ozone: this, coupled with the relatively high dosage rate required for fly ash treatment, can make this quite an expensive proposition.

Hurt et al identified the conditions for use of the gas to oxidize the carbonaceous material on some fly ash materials tested. To achieve the desired effect for foam index reduction, dosage ranges from 0.5 to 2 or 3 g of ozone/kg of fly ash. Ozone is toxic and needs to be utilized fully or broken down into atmospheric oxygen after the atomic oxygen has taken part in the reaction step. This in itself requires very careful management of the contacting and dosage rate or a back up catalytic breakdown system using manganese dioxide or thermal treatment to about 300° C. At the latter temperature, the residual ozone is reduced to negligible levels.

The authors also elaborated on the mechanism and noted that the actual LOI figure increased with the ozone application. This implies a different mechanism from a breakdown of carbonaceous material into components such as carbon dioxide and water vapor unless they are still held as by-products on the surface.

In international patent WO 02/097330 A1J.M, Tranquilla discloses the use of a microwave reactor together with a carbon-free material and oxygen contacting for reduction of the carbon content in high carbon fly ash. However, the operating temperatures employed with the technique are above 600° C., which leads to the expenditure of significant microwave energy for its attainment. This is, therefore, a variant on a high temperature process for burnout of carbon in fly ash. While this process reduces the carbon content significantly, it is not specifically targeted at lowering the foam index or ammonia removal. The low temperature and energy requirement is the stated objective of this present application.

Another form of energy that has been applied to accelerate reactions and, in particular, oxidations in the field of organic chemistry and wastewater treatment is ultraviolet radiation. However, this has insufficient energy, at close to ambient temperatures, to engage in burnout processes. It also requires relatively accessible surfaces, high surface area, thin layers of material, if the material is solid, or rapid material exchange within the body of the material to be effective.

Other inventors have sought to utilize chemical injection or spray treatment to modify the surface of the fly ash and passivate the fly ash surfactant demand. While this is a low temperature application, which minimizes the energy and is applied to dry fly ash, it has possible future unpredictable consequences for the concrete. Dosing and application rate are a practical issue, which are difficult to control with material that is being transferred at high rate into tankers for dispatch. Generally there is poor penetration into the heart of the flowing mass. The chemicals themselves are potentially hazardous if spilled in transit and are often aliphatic or aromatic carboxylic acids and their salts—see U.S. Pat. No. 6,599,358.

DISCLOSURE OF INVENTION

The present application seeks to beneficiate a variety of different coal burning power plant fly ash materials that either have a high foam index problem or are contaminated with ammonia or a combination of these issues and are not marketable into the cement/concrete industry. It also seeks to overcome the shortcomings of the aforementioned methods and provide a safe, economical method of treatment of ash.

In the methodology of the present application, a surface blocking mechanism is employed that minimizes the energy requirements for processing the ash. It does not require heating. The treatment only modifies superficial layers of the fly ash while the gaseous agent itself has a half-life that is measured in seconds or at most minutes. Fly ash is a commodity and cannot stand high costs in processing to bring it into a marketable state. Accordingly, what is proposed in this application is specifically a low cost method of upgrading the ash merely by localized surface treatment of the offending carbon. The unique aspect of the application is the careful administration of ionized air generated from ambient humid air for ionic treatment of the surface of the carbon utilizing a contacting method and environment operating at, or close to, ambient temperature. (Air is specifically mentioned due to its low cost, although oxygen or oxygen-enriched air may be used, provided there is sufficient humidity in it). Thus, the operational cost of heating material and the associated capital cost of thermal equipment is avoided.

An example of foam index treatment on a specific C-type fly ash is given below. The initial foam index was successfully reduced by ionized ambient air having a relative humidity of approximately 50% by the following

Method Dosage g/kg of fly ash Ionized 0.004 0.39 0.77 1.55 Air Out- Out- Input put Input put Input Output Input Output Foam 95 70  95 30 100 25 95 15 Index Reduction 26.3% 68.4% 75.0% 84.2% Ozone 0.31  0.61 1.22 3.06 Out- Out- Input put Input put Input Output Foam 95 85 105 80 105 90 95 80 Index Reduction 10.5% 23.8% 14.3% 15.7% amounts:

It should be noted that the target of foam index in this particular case is approximately 30. (In some instances, the measurements are made in milliliters rather than drops, as shown) However, the relative reduction is the indicator of the efficiency. For ionized air, the dosage rate reflects the equivalent ionic oxidizing power in g per kg of ash. Whereas with ozone it is the actual grams of O₃ passed through so many grams of sample-expressed as g/kg.

While there is some scatter in the results with dry ozone, it should be noted that on the same material and weight treated, the ozone tests did not achieve more than 24% reduction at a dose of 0.61 g/kg and never reached the desired reduction of around 70% even at much higher dosage rates up to 3.1 g/kg. By contrast, the ionized air reached the targeted value (30 drops) with only 0.39 g/kg-one eighth of the concentration of ozone, which in the highest dosage only reached 15.7% reduction (to 80 drops). Comparing the lightest dose of ionized air (0.004) against the heaviest of ozone (3.06) indicates the ability to exceed the performance of ozone on this material with over 700 times lower dosage.

The fly ash material needs to be tested to establish dosing rates and in certain cases dosage may be increased to treat material that has both foam index and high ammonia.

The disclosed system and method seeks to avoid a number of the issues noted with the above prior art in the following way:

Compared with thermal routes—

-   -   No fuel and much less overall energy is anticipated for the new         process     -   The system can be applied with relatively simple gas/solid         contactors without special construction requirements         Compared with the ozone route—     -   No expensive drying system to low dew points is needed     -   Some residual moisture level in the gas or the solid is an         advantage     -   Humid or ambient air may be utilized (or oxygen but only to         speed up the effect)     -   Dosage rates are one to two orders of magnitude less than with         ozone     -   The toxic excess is totally eliminated or greatly reduced     -   No expensive break down system or use of heat is required for         excess reactant     -   The system will work with both FI (foam index) problems and         ammonia     -   The final breakdown products are innocuous

Furthermore, if compared to some of the proposed options for introducing special surfactant-modifying chemicals, which incidentally have undergone no long term monitoring of their effect on resultant concrete properties, the technique leaves no registerable by-products or modifying chemicals. It has a short life in its effect and the by-product is oxygen. Hence, there is no deleterious effect on the concrete or cementitious properties of the ash when mixed with cement. In addition, as the reactant is administered in a gaseous form there is less risk of poor dosing rate or coverage leading to quality control issues.

-   -   With the present methodology, once the correct dose is         established from tests on the ash initially, the method is not         prone to the “hit and miss” syndrome with liquid injection or         spray methods of applying chemicals. These systems lead         potentially to downstream chemical component issues in the         concrete mix.

The ionized air can be generated through a device, which for example, has planar or concentric arrays of electrodes, without a dielectric intermediary to nullify the power arc or thermal discharge of the device. It does not require dried air or oxygen, which are needed for ozone—e.g. dew points of −40° C. for example. The presence of the moisture is beneficial in stabilizing the plasma gas that is generated. The electrical field creates ionic oxygen species and hydroxyl ions, which are highly reactive on suitable targets. These ions effectively block the surface of the active carbon sites. This ionic gas will not significantly react with massive carbon that is present from incomplete combustion burnout of the original coal particles. Hence, negligible change in loss on ignition is effected. Carbon burnout is not the objective.

The ionized gas will furthermore progressively attack adsorbed ammonia on sites on the surface of the carbon and mineral matter and complete the reaction of this to form innocuous nitrogen and water vapor. Hence, ionized air is capable of providing a solution to the oxidation and treatment of fly ash that is presently problematic and incapable of being sold due to either ammonia or foam index issues or both of these problems.

Other types of device including those with dielectric barriers and corona discharge or pulsed mechanisms can also generate ionized air. It is important that the excitation voltage and frequency, with the water vapor present, lead to ionized components, free radicals and hydroxyl ions, which take part rapidly in carbon surface reactions. Some of these are said to be at least two orders of magnitude more powerful than molecular ozone as reacting species.

The ionized air or ionized oxygen is not the low-level or background ionized air that is found frequently in domestic products for allergy or dust treatment. These devices have insufficient energy level to bring about the necessary reactions. This product is made from a high frequency wave. It can be sinusoidal but is preferably square, and creates an alternating electrical field that has 7-20 kV of peak voltage and a rise and fall time that exceeds 10⁶ volts/sec. The frequency and shape of the wave generator assure that the power arc cannot develop before the voltage potential is cut-off. The repeated excitation of the atoms produces a large number of ions in the cold plasma gas. While a dielectric may still be utilized in some designs, the manufacturing costs are minimized by eliminating the tolerance issues associated with ceramic tubes or quartz dielectrics, which must be made concentric in geometry with the outer and inner electrodes. Dielectric barriers only serve to diffuse the power and prevent arcing in a plasma reactor—creating a so-called low temperature corona discharge—about 700° K. or less.

A discussed previously, the presence of moisture or H₂O in the gas stream is actually beneficial. Many of the incoming H₂O molecules form hydroxyl ions or radicals inside the plasma reaction zone. Those that do not enter into reactions with other ions or break up serve to screen other ions. The H₂O molecule has an approximately 120-degree dipole, with partial charges on the two hydrogen atoms and the oxygen atom. These partial charges enable them to orient themselves as clusters around partially charged oxygen molecules and ions increasing their longevity. The gas is effectively stabilized until it contacts or is adsorbed onto the various carbonaceous film surfaces in the fly ash.

The dosing rate relative to fly ash will depend on the level of contamination and the particle size range—finer particles require higher dosage rates and certain types of fly ash are more intractable. As the aim is not to combust or react the carbon, provision of enough ions for coverage of the surface sites is the objective.

Within the scope of the present invention there are essentially three mechanisms; all operated at low temperature and all effectively surface oxidations that might be applied. In certain instances, to accommodate the variability or the intransigence of the contamination in the fly ash a combination of systems can be effective.

-   -   The fly ash from a given power plant site ideally needs to be         tested to determine the best sequence and level of energy for         the treatment process. Hence, it may require photolytic         breakdown with ultraviolet light, or microwave energy or ionized         air or some combination of all three. The common thread is that         the oxygen in the air is energized, largely without the         conventional application of heat for example in a combustion         process, leading to ionic formation and free radical reactions.         Thus, ionized air alone, ionized air with ultraviolet radiation         inside the contacting reactor to enhance the ionized air effect         and/or microwave radiation to accelerate the reaction on the         surface are all possible methods of enhancing the oxidation.         Again it is emphasized that other than local surface heating of         particles through reaction and radiant adsorption there is no         wholesale heating of the gas stream or bulk of the mineral         matter to combustion or near combustion temperatures. The         process is carried out at low temperatures or substantially the         mass of material is near or at ambient conditions. Some moisture         in the air or the natural relative humidity of the ambient air         is essential to the treatment process.

With both ultraviolet and microwave radiation, there is the need to contain these emissions within the contactor or reactor so that there is no harmful egress into the environment. However, the effect is localized and there are substantially no residual gases or chemicals that must be eliminated downstream.

Compared to ozone the power input required for the relevant amount of ionized air will be substantially less perhaps of the order of half of the power to make ozone and apply it to the fly ash. In addition, it might be expected that the capital cost of such equipment based on the principles indicated above will also be of the order of half of the ozone generator for similar duties.

Although it is possible to pass dilute phase solids in humid air through purposely designed plasma reactors and generate the ions in situ, the desired treatment effect is obtainable by first making the ionized gas stream and then contacting the fly ash particles.

The application of the ionize air or gas mixture to the fly ash is the next issue. Contact times and reactor geometries will be adapted from good engineering principles. These will include the ability to maximize the slip velocity or differential velocity of the particles relative to the gas stream—which in itself reduces the boundary layer effect and increases the overall mass transfer coefficient.

Suitable contacting devices range from pipeline or transfer line reactors, to fluidized beds, cyclonic reactors or especially toroidal fluidized beds as per U.S. Pat. Nos. 4,952,140 or 6,564,472, for example, (which have the high slip velocity mentioned earlier). In certain cases, the duty could be met with panel bed filter type configurations, packed and moving bed designs or even just baghouses adapted for the purpose. Depending on the level of contaminants, the application of ionized air may be made by injection into a silo or hopper containing the material. Here, the mixing and contacting may be poor but the residence time is extended. Contact times are a function of the device but can range from a few seconds to some minutes.

BRIEF DESCRIPTION OF DRAWINGS

The accompanying drawings illustrate preferred embodiments of the present invention according to the best mode presently devised for making and using the instant invention, and in which:

FIG. 1 is a flowchart of a preferred example of the disclosed invention.

FIG. 2 is a flow chart of another example of the inventive steps disclosed here.

FIG. 3 is yet another example of the inventive steps disclosed here, the process being carried out through a fluidized-bed reactor of the type sold under the Torbed trademark.

FIG. 4 is an example allowing for multiple reactors.

FIG. 5 illustrates a UV quartz reactor that may be used with the disclosed system to add exposure of ultra violet radiation to the fly ash.

FIG. 6 illustrates the use of ultraviolet radiation in a Torbed® type reactor.

BEST MODE FOR CARRYING OUT THE INVENTION

While the invention will be described and disclosed here in connection with certain preferred embodiments, the description is not intended to limit the invention to the specific embodiments shown and described here, but rather the invention is intended to cover all alternative embodiments and modifications that fall within the spirit and scope of the invention as defined by the claims included herein as well as any equivalents of the disclosed and claimed invention.

Turning now to the accompanying drawings, it will be understood that FIG. 1 indicates the conveyance of particulate fly ash 10 in a gas stream 12 from a feed hopper or silo 14, which contains the fly ash containing carbon to be treated, through a contactor or reactor 18 to a product hopper or silo 20. Generally, an ionized gas 22 can be an additive to the air stream that is conveying the fly ash. In certain cases, it may be appropriate to make all the ionized gas present in the conveying stream itself rather than by admixture. This is shown in FIG. 1 as the “or” case 24.

FIG. 2 shows the ionizer application with a fan delivering air through the energized zone 30 to the annular zone 32 of the reactor 18, carrying air and particles in at one end and out at the other. Although not shown here, it is also possible to design the ionizer with streamlined internals for actual passage of the solids in dilute phase through the reaction zone. In this case it is again important to have humidity in the transport air or gas so that the relevant species can be formed and interact heterogeneously with the fly ash surface. Hence, the plasma reactor itself and the contactor might be one and the same device, provided the solids are administered in a dilute or finely distributed phase.

FIG. 3 depicts a reactor for improving the contact time or mixing of the gas with the solids through the agency of a fluidized bed or a TORBED® reactor 40. (TORBED is the registered trademark of Mortimer Technology Holdings Ltd., UK). This method of contacting has low pressure drop and high mass transfer coefficient between gas and particle.

-   -   Either methodology has advantage where there is a need for         extended residence time.

In other instances, ionized air could be applied direct to a silo alone or in addition to a transferring reactor or contactor delivering to the silo. FIG. 4 shows the silo method of implementing the proposed method of treatment. This applies to situations where there is a need for even more residence time for contact. Two silos 32 are shown adapted for passage of ionized gas 34 from the bottom 36 upwards through the packed bed of ash 38. Ionized gas is introduced as ash is fed counter-currently into the silos.

-   -   The silos are cycled to treat material prior to discharge to         truck or rail car.

An experiment was carried out to determine if ultraviolet would effect ammonia breakdown reactions destroying ammonia compounds on fly ash. “Ultraviolet” covers a range of wavelengths ranging from short wave 254 nm to 312 nm, medium wave, to 365 nm, long wave, with the short wave being the most effective for rupturing of C—H bonds. Because N—H bonds have similar molecular bond energy it was thought that 254 nm wavelength UV might be effective at rupturing the bonds. The presence of humid air was thought to be advantageous due to the potential for formation of additional oxidizing species that are necessary for correction of foam index. The experiment therefore involved a sweep of humid air while the fly ash was irradiated. Being a surface reaction, an elongated geometry of reactor with shallow layer of fly ash was selected as shown in FIG. 5 below.

The mechanism for ultraviolet treatment is postulated to involve ammonia, as an adsorbed gaseous species only, and its breakdown into nitrogen and hydrogen due to the photolytic action:

2NH₃=N₂+2H₂

In the experiment, the uv light was operated intermittently on and off. During the off periods the fly ash was shaken to expose fresh material surface. With five periods of shaking, the sum of the “on” periods totaled 15 minutes and was therefore represented the total exposure time.

Exposure to ultraviolet light, UV-C at 254 nm, and 6 watts of power with 3 lpm of 50% RH airflow successfully produced a low ammonia level of 13.5 ppm in a C-ash having an untreated level of 121.5 ppm. It simultaneously had a foam index reduction from 95 to 75, (21%).

FIG. 6 depicts the in-situ application of ultraviolet radiation introduced down the center of a TORBED reactor or alternatively through uv-transparent windows embedded in the sidewalls, (as an example of a preferred embodiment). The reactor alternatively could have a microwave system with a wave-guide positioned internal to the reactor to achieve the same effect and may or may not have a separate external generating source of ionized air.

-   -   The diffuse cloud of particles that is generated inside this         type of reactor is ideal for the radiation and mass transfer.

Unlike ozone, no significant residual breakdown equipment for excess gas or ionized species is envisaged as the high surface area of particulates and the heterogeneous reactivity of the species is likely to utilize the majority of the gas. It is however possible to provide for the eventuality of a small amount of breakthrough with a fabric filter containing some activated carbon or even manganese dioxide—operated at ambient temperatures.

An objective of the present invention is to simplify the application and hence the cost of the system so system arrangements where the ionized air equipment becomes a simple add-on are a substantial benefit in limiting the overall cost of treating the fly ash.

Thus it can be appreciated that the above-described embodiments are illustrative of just a few of the numerous variations of arrangements of the disclosed elements used to carry out the disclosed invention. Moreover, while the invention has been particularly shown, described and illustrated in detail with reference to preferred embodiments and modifications thereof, it should be understood that the foregoing and other modifications are exemplary only, and that equivalent changes in form and detail may be made without departing from the true spirit and scope of the invention as claimed, except as precluded by the prior art. 

1. A method for treating carbon-containing fly ash to reduce the adsorption capacity of the contained carbon, the method comprising: providing a gas stream containing ionized air; providing an amount of fly ash containing carbon having an adsorption capacity; exposing the fly ash to the gas stream to expose the carbon to the ionized air to reduce the adsorption capacity of the carbon.
 2. The method of claim 1 wherein said ionized air is produced by exposing a stream of air to an alternating electrical field having a peak voltage of seven to twenty kV of peak voltage and a voltage rise and fall that exceeds 10⁶ volts per second.
 3. The method of claim 2 wherein said air has a high relative humidity, and said fly ash contains ammonia, so that the ammonia and water react with the fly ash to create an oxidizing species that further reduces the adsorption capacity of the carbon.
 4. The method of claim 3, wherein said gas stream containing ionized air is at a temperature below that required for oxidation of substantial amounts of the carbon.
 5. The method of claim 4 and further comprising exposing the fly ash to ultraviolet light.
 6. The method of claim 5 wherein said ultraviolet light comprises UV-C at 254 nm. 